Stockholm Convention on Persistent Organic Pollutants
Persistent Organic Pollutants Review Committee
(POPRC)
DRAFT RISK PROFILE
For
Commercial Octabromodiphenyl Ether
Draft prepared by:
The ad hoc working group on commercial octabromodiphenyl ether
May, 2007
1
Draft Risk Profile for Commercial Octabromodiphenyl Ether
Note:
In accordance with the procedure laid down in Article 8 of the Stockholm
Convention, this draft was prepared by the Persistent Organic Pollutants Review
Committee (POPRC) during its inter-sessional work. Parties and observers to the
Stockholm Convention are invited to provide technical and substantive comments on
this draft. Comments received will be considered by the ad hoc working group and the
revised draft will be made available for the third meeting of the POPRC (19-23
November in Geneva). Please submit your comments to the Secretariat of the
Stockholm Convention preferably by e-mail before July 1, 2007 to:
Secretariat of the Stockholm Convention
POPs Review Committee
11-13 chemin des Anémones
CH-1219, Châtelaine, Geneva, Switzerland
Fax: (+41 22) 917 80 98
E-mail: ssc@pops.int
___________________________________________________________________________________
Ad hoc working group on commercial octabromodiphenyl ether
Chair:
Ms. Jacqueline Alvarez (Uruguay)
Drafter: Mr. José Tarazona (Spain)
Members: Mr. Ian Rae (Australia), Mr. Robert Chénier (Canada), Mr. Jianxin Hu
(China), Ms. Liselott Säll (Norway), Ms. Evlin Fabjan (Slovenia), Mr. Bo
Wahlström (Sweden), Ms. Leena Ylä-Mononen (designated by the United
Kingdom), Mr. Al El-Shekeil (Yemen)
Observers:
Mr. Lee Eeles (Australia), Mr. Lars Juergensen (Canada), Mr. Wenchao
Zang (China), Mr. Timo Seppäla (Finland), Ms. Sandrine Andres (France),
Ms. Indrani Chandrasekharan (India), Mr. Takashi Fukushima (Japan), Mr.
Dzierzanouski (Poland), Ms. Bettina Hitzfeld (Switzerland), Ms. Sekai
Ngarize (United Kingdom), Mr. Chris Blunck (USA), Mr. Robert Campbell
(USA), Mr. Alan Rush (USA), Mr. Kenneth Moss (USA), Mr. Sylvain
Bintein (EC), Mr. Masayoshi Shibatsuji (WHO), Mr. Joseph DiGangi (EHF),
Mr. Mark Trewhitt (CropLife Int.)
___________________________________________________________________________________
This draft risk profile is prepared on behalf of the European Union and its Member
States by Dr José V. Tarazona, Director of the Department of the Environment of INIA,
Spain in cooperation with Dr E. Alonso, Dr. MA Martinez, A de la Torre and P Sanz,
Environmental Department, CIEMAT, Spain and the Spanish National Reference
Centre for POPs for the European Commission, DG Environment.
2
Table of Contents
EXECUTIVE SUMMARY .............................................................................................. 4
1. INTRODUCTION ........................................................................................................ 6
1.1 Chemical identity of the proposed substance ..................................................... 6
1.2 Conclusion of the POP Review Committee of Annex D information ................ 8
1.2.1.
Persistence .............................................................................................. 11
1.2.2.
Bioaccumulation ..................................................................................... 11
1.2.3.
Potential for long-range environmental transport ................................. 12
1.2.4.
Adverse effects ........................................................................................ 12
1.2.5.
Statement of the reasons for concern ..................................................... 13
1.3 Data sources .......................................................................................................... 13
1.4 Status of the chemical under international conventions ....................................... 14
2 SUMMARY INFORMATION RELEVANT FOR THE RISK PROFILE ................ 14
2.1 Sources ................................................................................................................. 14
2.2 Environmental fate ............................................................................................... 15
2.2.1 Persistence ..................................................................................................... 15
2.2.2 Bioaccumulation ............................................................................................ 16
2.2.3 Long range environmental transport ............................................................. 17
2.3 Exposure ............................................................................................................... 18
2.3.1 Atmosphere.................................................................................................... 18
2.3.2 Water ............................................................................................................. 18
2.3.3 Sediments ...................................................................................................... 18
2.3.4 Soil ................................................................................................................. 19
2.3.5 Waste Effluent and Biosolids ........................................................................ 19
2.3.6 Biota .............................................................................................................. 19
2.3.7 Humans .......................................................................................................... 21
2.4 Hazard assessment for endpoints of concern ........................................................ 22
3 SYNTHESIS OF THE INFORMATION .................................................................... 25
4 CONCLUDING STATEMENT .................................................................................. 27
EXECUTIVE SUMMARY
The European Union and its Member States, which are Parties to the Stockholm
Convention, submitted a proposal in July 2006 for listing octabromodiphenyl ether in
Annex A of the Stockholm Convention pursuant to paragraph 1 of Article 8 of the
Convention, and the POPRC agreed that the commercial product Commercial
octabromodiphenyl ether – actually a mixture as described below - met the screening
criteria of Annex D to the Convention. This risk profile reviews the available information
on the commercial mixture and its main components: Hexa, Hepta, Octa and
NonaBDE.
The polybrominated diphenyl ethers in general are used as flame retardants of the
additive type. They are physically combined with the material being treated rather than
chemically combined (as in reactive flame retardants). The commercial products cover
several congeners and bromination levels. The information provided by the bromine
industry indicates that the octa commercial product has been produced in The
Netherlands, France, USA, Japan, UK and Israel, but since 2004, it is no longer
produced in the EU, USA and the Pacific Rim and there is no information that indicates
it is being produced in developing countries. According to the Bromine Science and
Environmental Forum (BSEF), OctaBDE was commercialized sometime in the mid
70’s. By the early 2000’s global production was <4000 tonnes/year and by the time
production ceased, demand was <500 tonnes; assuming 30 years of production at
6000 tonnes per year total production volume would be around 180,000 tonnes.
Assuming that the commercial octaBDE is not longer produced, the releases to the
environment must be associated to historical processes, as well as to releases during
the service life of articles containing the commercial mixtures and at the end of article
service life during disposal operations. Switzerland reported for this country diffuse
emission from the use of products containing OctaBDE of about 0.37 t/a (based on
worst-case estimations) for a total stock of 680 tons.
The persistence of these PBDE in the environment is well documented. The only
relevant degradation pathways identified until now are photolysis, anaerobic
degradation and metabolism in biota, acting through debromination and producing
other BDE which may have higher toxicity and bioaccumulation potential.
The bioaccumulation potential for sediment exposure and particularly for exposure via
food is well documented for some c-OctaBDE components. There is also enough
toxicokinetic information demonstrating that elimination rates in some vertebrate and
invertebrate species are equivalent to those observed for other POPs, with values in
the range of 0.01 to 0.5 days-1, equivalent to a half life of about 14 to 70 days
assuming first order kinetic. Thus a bioaccumulation potential is confirmed at least for
some isomers, as well as biomagnification in some food chains. As debromination into
other POP-like chemicals is suggested to be a relevant contribution to the dissipation of
hexa to nonaBDE, the absence of food-chain biomagnification for a specific congener
on a specific taxonomic group does not necessarily decrease the overall concern.
In fact, biota monitoring data in remote areas offer the best demonstration on the
potential for long range transport of c-OctaBDE components, in particular for Hexa and
HeptaBDE. Theoretically this presence could also be explained by the transport of
DecaBDE and its subsequent debromination. However, the comparative analysis of the
available information on the physical-chemical properties of the different PBDE
homologues indicates that debromination from DecaBDE might contribute to the
process but it is not realistic to assume that this explains the process without additional
4
transport from other congeners. Thus, based on the available information a long-range
transport is expected for the c-OctaBDE components, and the role of atmospheric
transport is confirmed at least for Hexa and HeptaBDE based on its detection in alpine
lakes.
Unfortunately, the available information on the toxicity and ecotoxicity of hexa to
nonaBDE is very limited and does not offer enough information for presenting sound
toxicological and ecotoxicological profiles for each isomer, mixtures of isomers and
commercial mixtures.
No relevant effects have been observed in aquatic, sediment and soil laboratory
studies. However, the measured endpoints and the exposure conditions employed in
some assays may be insufficient for a proper assessment of chemicals such as hexa
to nonaBDE.
The available information on mammals and birds offer relevant information. The lowest
reported NOAEL for traditional endpoints is 2-5 mg/kg bw/d. The effects are relevant
for the health and the ecological assessments and therefore useful for assessing risks
for humans and wildlife. In addition, immuno-toxicological effects and particularly
developmental neurotoxic effects observed after a single dose require specific
attention. A critical body burden for hexa BDE 153 of 2000 µg/kg lipid has been
estimated based on a NOEL of 0.45 mg/kg; it should be noted that hexa BDE 153
concentrations close to this value have been found in several species and geographic
sites and total PBDE concentrations frequently exceed largely this threshold.
The evaluation of the human and environmental risk of commercial OctaBDE
associated to its potential for long range transport is not an easy task as the
commercial product is a mixture of components with different properties and profiles,
which may also be released to the environment due to its presence as components of
other PBDE commercial products and also produced in the environment by
debromination of commercial decaBDE.
The greatest difficulty appears for the estimation of the potential hazard of the
commercial mixture and its components. There are traditional ecotoxicological and
toxicological studies where no effects have been observed even at unrealistically high
concentrations. However, an in-depth assessment of these studies considering in
particular the properties and toxicokinetic of PBDE indicates that the test design,
exposure conditions and measured endpoints are not appropriate for a sound
assessment of these types of chemicals. Thus, the lack of effects reported in those
tests should be considered with care.
In addition, specific studies have reported particular hazards such as delayed
neurotoxicity and immunotoxicity which may be particularly relevant in the assessment
of both human health and ecosystem risks.
Based on the existing evidence, additional concerns related to the debromination into
toxic BDEs, the increasing evidence relating these chemicals with other POPs
(similarities between PBDEs and PCBs; relationships with dioxins and furans), and that
under Article 8, paragraph 7(a) of the Convention the lack of full scientific certainty shall
not prevent a proposal from proceeding, it is concluded that the components of cOctaBDE, Hexa to NonaBDE, are likely, as a result of LRET, to lead to significant
adverse human health and/or environmental effects, such that global action is
warranted.
5
1. INTRODUCTION
The Stockholm Convention is a global treaty to protect human health and the
environment from persistent organic pollutants (POPs), of which twelve are currently
listed under the Convention. POPs are chemicals that remain intact in the environment
for long periods, become widely distributed geographically, accumulate in living
organisms and can cause harm to humans and the environment. The European Union
and its Member States, which are Parties to the Stockholm Convention, submitted a
proposal in July 2006 for listing octabromodiphenyl ether in Annex A of the Stockholm
Convention pursuant to paragraph 1 of Article 8 of the Convention, and the POPRC
agreed that the commercial product Commercial octabromodiphenyl ether – actually a
mixture as described below - met the screening criteria of Annex D to the Convention.
1.1 Chemical identity of the proposed substance
This proposal concerns the c-OctaBDE. There are several components in the
commercial product, with different properties and potential risks. Thus this risk profile
focuses on the assessment of individual components of the commercial product, and
the final compilation for an overall assessment of the commercial product itself.
It is believed that little if any c-OctaBDE is produced since the major supplier located in
North America stopped production in 2004. The commercially supplied OctaBDE was
complex mixture consisting (as of 2001 within the EU Member States) typically of
≤0.5% Pentabromodiphenyl ether isomers, ≤12% Hexabromodiphenyl ether isomers,
≤45% Heptabromodiphenyl ether isomers, ≤33% OctaBDE isomers, ≤10%
Nonabromodiphenyl ether isomers and ≤0.7% Decabromodiphenyl ether. The
composition of older products or products from non-EU countries may be different from
this.
The c-OctaBDE is sold as a technical grade under the Chemical Abstracts Service
(CAS) Registry number for the OctaBDE isomer.
IUPAC Name:
Diphenyl ether, octabromo derivative (octabromodiphenyl ether,
OctaBDE)
Synonyms: octabromobiphenyl oxide, octabromodiphenyl oxide, octabromo
phenoxybenzene and benzene, 1,1’ oxybis-, octabromo derivative
CAS Number:
32536-52-0
Molecular formula: C12H2Br8O
Molecular weight:
801.38
Chemical structure:
Three polybrominated diphenyl ether flame retardants were historically available
commercially. They are referred to as penta, octa and decabromodiphenyl ether, but
each product is a mixture of diphenyl ethers with varying degrees of bromination.
6
Several synonyms and abbreviations for polybrominated diphenyl ethers exist and
these are shown below:
polybrominated biphenyl ethers ≡ polybromobiphenyl ethers – PBBEs
polybrominated biphenyl oxides ≡ polybromobiphenyl oxides - PBBOs
polybrominated diphenyl ethers ≡ polybromodiphenyl ethers - PBDPEs
polybrominated diphenyl oxides ≡ polybromodiphenyl oxides – PBDPOs
The compositions of the commercial polybrominated diphenyl ethers based on
composite samples from the EU suppliers are shown in Table 1. These are the
substances that have been used in the recent tests and used as a basis for the EU risk
assessment reports for the three commercial substances. These data indicate that if
tetra- and pentabromodiphenyl ethers are present in the commercial
octabromodiphenyl ether or Decabromodiphenyl ether products, they must be present
only at very low levels.
Table 1. Composition of commercial polybrominated diphenyl ethers as described in
the EU RAR.
There is some discrepancy between the composition of octabromodiphenyl ether given
in the OECD Voluntary Industry Commitment (VIC) and the composition more recently
supplied (Table 1), particularly with regard to the levels of the pentabromodiphenyl
ether congener. The composition given in the VIC is as follows:
Hexa/pentabromodiphenyl ether 1.4-12.0%1
Heptabromodiphenyl ether 43.0-58.0%
Octabromodiphenyl ether 26.0-35.0%
Nonabromodiphenyl ether 8.0-14.0%
Decabromodiphenyl ether 0.0-3.0%
In the VIC it is not clear how much if any pentabromodiphenyl ether is actually present.
No details of the analyses used were provided. Also, at the time the VIC was set up,
production of octabromodiphenyl ether was carried out in the EU. Since then,
production moved to sites outside the EU, and some producers have stopped
producing octabromodiphenyl ether altogether. This may have had some effect on the
composition. From the information presented in Table 1 above, it is clear that if
1
The Bromine Science and Environmental Forum (BSEF) suggest that the discrepancies are related to
analytical limitations at the time, this represents a total of PentaBDE and HexaBDE congeners, however
the majority of this % is believed by BSEF to be the hexaBDE fraction.
7
pentabromodiphenyl ether is present in the commercial product, it will be at much lower
levels than the 12% indicated by the VIC. La Guardia et al (2006) have recently
reported additional information on the composition of commercial mixtures.
The commercial mixture covered by this entry is therefore a complex combination of
isomers and congeners, as defined at POPRC.
There is a tendency in scientific literature to present the identities of polybrominated
diphenyl ether congeners using the numbering system based on the polychlorinated
biphenyl system. This risk profile will focus on the series of hexa, hepta, octa and nona
homologues:




Hexabromodiphenyl ethers (benzene, 1,1'-oxybis-, hexabromo derivative;
hexaBDE) (CAS No. 36483-60-0; IUPAC Nº between BDE-128 and BDE-169)
Heptabromodiphenyl ethers (benzene, 1,1'-oxybis-, heptabromo derivative;
heptaBDE) (CAS No. 68928-80-3; IUPAC Nº between BDE-170 and BDE-193)
octabromodiphenyl ethers (benzene, 1,1'-oxybis-, octabromo derivative;
octaBDE) (CAS No. 32536-52-0; IUPAC Nº between BDE-194 and BDE-205)
Nonabromodiphenyl ethers (benzene, 1,1'-oxybis-, nonabromo derivative;
nonaBDE) (CAS No. 63936-56-1; IUPAC Nº between BDE-206 and BDE-208)
The complexity for setting a risk profile for a complex mixture has been already
discussed by the POPRC with reference to the commercial mixture of
pentabromodiphenyl ether, and the situation is similar for the commercial mixture of
octabromodiphenyl ether. Briefly, there are three main conceptual issues:



Each isomer and congener may have different physicochemical properties,
persistence, bioaccumulation potential, toxicological and ecotoxicological
profiles and potential for long range transport
All, most or several isomers and congeners in the mixture may act through the
same mechanism of action and the assessment of the individual risk profiles
may not be enough for a proper estimation of the overall risk of the commercial
mixture due to additive and synergistic effects.
The debromination in the environment and biota represents an additional
potential source of bromodiphenyl ethers and related metabolites. The
metabolites may be more bioavailable and/or toxic than the parent compounds.
The current complexity when analysing this situation is increased by the reduced
availability of information as the physical-chemical, fate, and (eco)toxicological
information covers in some cases assays with the commercial mixtures, while in other
cases the studies focused on mixtures of isomers and/or homologues, or individual
compounds. A full data set for conducting a risk profile is not available for the
commercial mixture or for the individual components. Thus the available pieces of
information have been combined in this risk profile. The report will present whenever
possible the risk expected for the commercial mixture.
1.2 Conclusion of the POP Review Committee of Annex D information
POP RC has evaluated Annex D information and has concluded that proposal fulfils the
requirements of Article 8 and Annex D of the Convention. The POPRC decision is
included below:
8
Annex to decision POPRC-2/6
Evaluation of commercial octabromodiphenyl ether against the
criteria of Annex D
A.
Background
1.
The primary source of information for the preparation of this evaluation was the
proposal submitted by the European Community and its member States that are Parties to
the Convention, contained in document UNEP/POPS/POPRC.2/INF/4.
2.
Additional sources of scientific information included critical reviews prepared by
recognized authorities, including the European Union risk assessment report on diphenyl
ether, octabromo derivative.
B.
Evaluation
3.
The proposal was evaluated in the light of the requirements of Annex D, regarding
the identification of the chemical (paragraph 1 (a)) and the screening criteria (paragraphs
1 (b)–(e)):
(a)
Chemical identity:
(i)
Adequate information was provided in the proposal and supporting
information. The proposal relates to commercial
octabromodiphenyl ether;
(ii)
The chemical structure for the pure compound octabromodiphenyl
ether was provided. Commercial octabromodiphenyl ether is a
mixture of several polybrominated diphenyl ethers and congeners
(pentabromodiphenyl ether isomers, hexabromodiphenyl ether
isomers, heptabromodiphenyl ether isomers, octabromodiphenyl
ether isomers, nonabromodiphenyl ether isomers and
decabromodiphenyl ether isomers);
The chemical identity of commercial octabromodiphenyl ether and the pure
compound octabromodiphenyl ether is adequately established;
(b)
Persistence:
(i)
There was no degradation in an OECD test (301D) over 28 days
(Ref. 3);
(ii)
Elevated concentrations of polybromodiphenyl ethers, including
octa and hepta bromodiphenyl ether congeners, were found in
agricultural soil more than 20 years after treatment of the soil with
contaminated sewage sludge, which is consistent with very long
half-lives for components of commercial octabromodiphenyl ether
(Ref. 2);
There is sufficient evidence that commercial octabromodiphenyl ether meets the
persistence criterion;
(c)
Bioaccumulation:
(i)
The log Kow value for the commercial product has been determined
to be around 6.29 (Ref. 3). Experimental results presented in the
European Union risk assessment report indicates that octa and
heptabromodiphenyl ethers have low bioconcentration factors (less
than 10–36); these results have been confirmed by data presented
and peer reviewed by the Japanese Government. Nevertheless, other
brominated diphenyl ethers present in commercial
octabromodiphenyl ether have been found to have higher
bioconcentration factors, for example 11,700–17,700 for
pentabromodiphenyl ethers (Ref. 3) and 1,000–5,600 for
hexabromodiphenyl ethers (Ref. 3);
9
(ii) and (iii) Field data provide evidence for the potential for
bioaccumulation of heptabromodiphenyl ether. Concentrations of
220–270 ng/g lipid weight in eggs of the peregrine falcon in
northern Sweden and Greenland have been reported (Refs. 4 and 5).
This evidence demonstrates that, despite its large molecular weight,
the molecule is found in top predators at levels similar to those of
bioaccumulable tetra and penta bromodiphenyl ether. In addition,
the estimated half-life in humans is 100 days (Ref. 6), suggesting a
potential for bioaccumulation. In soil biota, the soil organism
accumulation factor for octabromodiphenyl ether 197 has been
calculated as 2 (Ref. 2).
There is sufficient evidence that commercial octabromodiphenyl ether meets the
bioaccumulation criterion;
(d)
Potential for long-range environmental transport:
(i) and (iii) The vapour pressure of commercial octabromodiphenyl ether is
reported to be 6.59 x 10-6 Pa at 21°C (Refs. 1 and 3). The
atmospheric half-life of the pure compound octabromodiphenyl
ether is estimated to be 76 days, which means that long-range
transport is possible for the substance;
(ii)
Monitoring data show that the hexa and hepta bromodiphenyl ether
congeners are present in biota in remote regions (Refs. 7 and 8) and
in Arctic air (Ref. 9);
There is sufficient evidence that commercial octabromodiphenyl ether meets the
criterion on potential for long-range environmental transport;
(e)
Adverse effects:
(i)
There are no data provided on the direct toxicological effects of
commercial octabromodiphenyl ether or polybromodiphenyl ether
congeners in humans;
(ii)
There is evidence of reproductive toxicity in mammals. The lowest
no observed adverse effect level (NOAEL) from the available
mammalian toxicity data for the commercial octabromodiphenyl
ether product was determined as 2 mg/kg bw/day in a
developmental study in rabbits (Ref. 3). Additional information on
the developmental toxicity of octabromodiphenyl ether has been
published recently (Ref. 10);
There is sufficient evidence that commercial octabromodiphenyl ether meets the
criterion on adverse effects;
C.
Conclusion
4.
The Committee concluded that commercial octabromodiphenyl ether meets the
screening criteria specified in Annex D.
The
bases for
this
conclusion
were
presented
in the document
UNEP/POPS/POPRC.2/12 – Summary of octabromodiphenyl ether proposal. The key
parts of this document, relevant for this risk profile, are reproduced below under
paragraphs 1.2.1 to 1.2.5, please note that text included here is the text from the
mentioned document ant that the discussion at POPRC2 focused on the fulfilment of
Annex D criteria and therefore did not covered all these issues.
10
1.2.1.
Persistence
OctaBDE has been found to photodegrade rapidly in a mixture of organic solvents, with a half-life
of around 5 hours, but the environmental significance of such a finding is uncertain (European
Commission, 2003). Besides, octaBDE is predicted to adsorb strongly onto sediment and soil,
which means that only a fraction of this PBDE will be exposed to sunlight, thus having the
potential to photodegrade. No information is available on the hydrolysis of octaBDE, but it is not
expected to be an important process for octaBDE in the environment.
Regarding biotic degradation, octaBDE is not readily biodegradable in standard tests (no
degradation seen over 28 days) and is not expected (by analogy with other brominated diphenyl
ethers) to degrade rapidly under anaerobic conditions. Nevertheless, other more highly
brominated congeners (deca and nonabromodiphenyl ether) have been found to degrade
anaerobically in sewage sludge, although at a very slow rate (Gerecke et al. 2005). The evidence
seems to indicate that there is little significant biotic or abiotic degradation of octaBDE.
It's worth noting that degradation of polybrominated diphenyl ethers (PBDEs) can yield
byproducts that are lower brominated congeners. For instance, Ahn et al. (2006) showed that
decaBDE immobilised on specific soil/sediment and mineral aerosols yielded a number of penta
to triBDEs, via octaBDE as an intermediate step. This may pose an additional environmental
concern, as these lower brominated diphenyl ethers are usually more toxic and much more
bioaccumulative.
1.2.2.
Bioaccumulation
The log octanol-water partition coefficient (log Kow) value for the commercial product has been
determined to be around 6.29 (European Commission, 2003). Based on its log Kow, octaBDE
congener would be expected to be bioaccumulative. However, the experimental result indicates
that octaBDE does not bioconcentrate (BCF<9.5), probably due to its large size, which may
preclude the crossing of cell walls in organisms.
Nevertheless, other brominated diphenyls present in c-octaBDE have been found to have higher
BCFs, for example:
11 700 – 17 700 for pentaBDE (European Commission, 2003); up to 5 600 for hexaBDE
(European Commission, 2003).
Thus, lower brominated diphenyls have BCF that meet perfectly the accumulation criteria. As
they are not only present in c-octaBDE (penta and hexaBDE make up to 12% of the commercial
product) but may also appear as a result of the degradation of the higher brominated diphenyls,
c-octaBDE can be considered to be bioaccumulative.
The EU Risk Assessment Report (European Commission, 2003) reports that brominated diphenyl
ethers with bromine contents both lower and higher than octaBDE have been detected in some
biota samples, notably predatory birds’ eggs. Theoretically, higher brominated congeners
shouldn't accumulate, as they are large molecules which are not likely to go through cell walls.
However, the work of Sellström et al. (2005) shows a noticeable accumulation of these
substances (hepta and decaBDE, amongst other BDEs) in wild falcons. Verreault et al. (2005)
found accumulation of several octaBDE congeners (both higher and lower brominated) in several
environmental samples of two Arctic top predators, and De Wit et al. (2006) reported a variety of
PBDEs in the Arctic. Therefore, a similar behaviour could be expected from octaBDE. In addition,
other studies (Tomy et al. 2004, Stapleton et al. 2004) mention that biotransformation of PBDEs
via debromination can lead to bio-accumulation parameters higher than expected, and a
consequent biomagnification risk.
By using the benchmark approach proposed by Scheringer (1997) and Beyer et al. (2000) (which
suggests that the intrinsic properties of a substance may be evaluated by studying those of
similar substances for which more data exist), it is likely that octaBDE is bioaccumlative.
11
1.2.3.
Potential for long-range environmental transport
In the EU Risk Assessment Report (European Commission 2003), the vapour pressure of
c-octaBDE is reported to be 6.59 x10-6 Pa at 21 °C. Brominated diphenyl ethers as a group all
have low vapour pressures, the vapour pressure tending to decrease with increasing bromination.
In the same report, the atmospheric half-life for octaBDE is estimated to be 76 days which means
that long-range transport is possible for this substance.
Table 1: Water solubility (WS), vapour pressure (VP) and Henry’s Law Constant (HLC) (at 25 °C)
for c-octaBDE and currently listed POPs
Substance
c-octaBDE *
WS mg/L
VP Pa
HLC Pa m3/mol
0.0005
6.59 x 10-6
10.6
POP-min
0.0012 (DDT)
2.5 x 10-5 (DDT)
0.04 (endrin)
POP-max
3.0 (toxaphene)
27 (toxaphene)
3726 (toxaphene)
0.5 (dieldrin)
0.04 (heptachlor)
267 (heptachlor)
POP-2nd max
* EU Risk Assessment Report
Table 1 shows the water solubility, vapour pressure and Henry's law constant for c-octaBDE, in
comparison with the maximum and the minimum for currently listed POPs. Henry's law constant,
a key property to determine if there is risk of long-range environmental transport for a substance,
is well inside the range set by the other POPs. Considering this fact together with its half-life, it
can be concluded that c-octaBDE is quite likely to undergo long-range environmental transport.
There are no monitoring data from remote locations available for octaBDE itself. In general,
PBDE concentrations have increased exponentially in arctic biota over the past two decades. The
lower brominated congeners (e.g. pentabromodiphenyl ethers and hexabromodiphenyl ethers)
present in c-octaBDE appear to be subject to long-range environmental transport, possibly via the
atmosphere, as they are widely found in sediment and biota in remote areas (Environment
Canada, 2004).
For other brominated congeners, hepta and decaBDE have been demonstrated to occur in
airborne particles in the high arctic (Wang et al., 2005). The modelling study by Wania and
Dugani (2003, as reviewed in European Commission 2004) concluded that decabromodiphenyl
ether was likely to be almost exclusively adsorbed to atmospheric particulates that would
effectively control the long-range transport behaviour of the substance. Besides, the presence of
decaBDE in moss in relatively remote regions of Norway, and in birds and mammals in Polar
Regions, has been attributed to long-range particulate transport (European Commission, 2004).
In summary, the data available for lower and higher brominated congeners (some of them also
present in c-octaBDE) show that they have potential for long-range environmental transport.
Analysis of c-octaBDE's chemical properties seems to support this conclusion, as Henry's law
constant is very similar to those of acknowledged POPs. Therefore, it can be expected that coctaBDE is subject to long-range environmental transport.
1.2.4.
Adverse effects
The available ecotoxicity data for the c-octaBDE product show little or no effect on aquatic
organisms (short-term fish study and a longer-term Daphnia magna study), sediment organisms
(Lumbriculus variegatus) and soil organisms (three species of plant and earthworms Eisenia
fetida) (European Commission 2003). However, the EU Risk Assessment Report identifies a risk
of secondary poisoning in other species (via ingestion of earthworms) for the hexabromodiphenyl
ether component in the c-octaBDE product (from use in polymer applications).
12
The EU Risk Assessment Report (European Commission 2003) reviews the available
toxicological studies on octaBDE. In that report, the lowest no observed adverse effect level
(NOAEL) from the available mammalian toxicity data for the c-octaBDE product is determined as
2 mg/kg bw/day in a developmental study with rabbits. Using this data, a predicted no-effect
concentration (PNEC) of 6.7 mg/kg food was derived in the EU Risk Assessment Report. Within
the EU, c-octaBDE has been classified as “Toxic”, due to its effects on human health, with the
risk phrases "may cause harm to unborn child", and "possible risk of impaired fertility".
The presence of lower brominated diphenyl ethers in the c-octaBDE products is of concern also
from the human health point of view as they are likely to have a higher potential to cause adverse
effects. WHO (1994) and more recently Birnbaum and Staskal (2004) have reviewed the
toxicological data on PBDEs in general.
All the abovementioned studies and assessments provide evidence that c-octaBDE causes
adverse effects. The possible formation of brominated dibenzo-p-dioxins and dibenzofurans
during combustion or other high temperature processes involving articles containing c-octaBDE is
another cause of concern (European Commission, 2003).
1.2.5.
Statement of the reasons for concern
The proposal of the European Union and its member States contains the following statement of
concern:
“The fact that c-octaBDE consists of several polybrominated diphenyl ethers and congeners
makes the assessment of POP characteristics more difficult than in the case of a single
compound. However, it can be concluded that c-octaBDE meets the criteria for persistence,
potential for long range environmental transport and potential to cause adverse effects. The
situation with regards to the screening criteria for bioaccumulation is not so clear cut but the
commercial product does contain at least a component group that has been confirmed by the
POPRC to meet all the screening criteria (pentabromodiphenyl ether). It also contains hexaBDE,
another congener with POP characteristics.
A second aspect of concern is that although the higher brominated BPDEs are
persistent, there is evidence that they can degrade under some conditions. Lower brominated
diphenyl ether congeners have been identified among the degradation products. Since some of
the products may be more bioaccumulative and toxic than the parent compound, any significant
formation would be a cause for concern.
An additional risk is the possible formation of brominated dibenzo-p-dioxins and dibenzofurans
during combustion and other high temperature processes involving articles treated with coctaBDE flame retardants.
Marketing and use of octaBDE has been prohibited recently in the EU but it is assumed still to be
produced and used as a flame retardant in many countries. As octaBDE and its congeners can
move far from their sources, single countries or groups of countries alone cannot abate the
pollution caused by it. Due to the harmful POP properties and risks related to its possible
continuing production and use, international action is warranted to eliminate this pollution.”
1.3 Data sources
The EU risk assessment report (European Commission 2003), the Canadian
assessment (Environment Canada, 2004), and references from the WHO (1994) report
were the main source of information used by the POP RC in Annex D screening.
Additional information has been submitted by Canada, the Czech Republic, Germany,
Lithuania, Norway, Switzerland, Turkey, UK, USA, the NGO Environmental Health
Fund on behalf of the International POPs Elimination Network (IPEN), and the industry
organization Bromine Science and Environmental Forum. Considering the large
13
amount of new scientific information produced nowadays, a review of recent scientific
literature has also been conducted and used as an essential data source in this report.

Note: additional information to be incorporated as a separate POP RC INF
document)
1.4 Status of the chemical under international conventions


OSPAR Convention: Octa-BDE takes part of the list of selected substances for
the OSPAR lists (no 236). Under the reviewed list, Octa-BDE is put under
section C – about the substances put on hold because they are not produced
and/or used in the OSPAR catchment or are used in sufficiently contained
systems making a threat to the marine environment unlikely.
UNECE, Convention on Long-range Transboundary Air Pollution (LRTAP) and
its Protocol on Persistent Organic Pollutants (POPs): c-OctaBDE is being
considered under Protocol procedures for inclusion.
2 SUMMARY INFORMATION RELEVANT FOR THE RISK
PROFILE
2.1 Sources
The information provided by the bromide industry indicates that the commercial product
has been produced in The Netherlands, France, USA, Japan, UK and Israel, but since
2004, it is no longer produced in the EU, USA and the Pacific Rim and there is no
information that indicates it is being produced in developing countries.
The polybrominated diphenyl ethers in general are used as flame retardants of the
additive type. They are physically combined with the material being treated rather than
chemically combined (as in reactive flame retardants). This means that there is the
possibility that the flame retardant may diffuse out of the treated material to some
extent.
Industry indicates that octabromodiphenyl ether is always used in conjunction with
antimony trioxide. In Europe, it is primarily used in acrylonitrile-butadiene-styrene
(ABS) polymers at 12-18% weight loadings in the final product. Around 95% of the total
octabromodiphenyl ether supplied in the EU is used in ABS. Other minor uses,
accounting for the remaining 5% use, include high impact polystyrene (HIPS),
polybutylene terephthalate (PBT) and polyamide polymers, at typical loadings of 1215% weight in the final product. In some applications, the flame retardant is
compounded with the polymer to produce pellets (masterbatch) with slightly higher
loadings of flame retardant. These are then used in the polymer processing step to
produce products with similar loadings as given above.
The flame retarded polymer products are typically used for the housings of office
equipment and business machines. Other uses that have been reported for
octabromodiphenyl ether include nylon and low density polyethylene (WHO, 1994),
polycarbonate, phenol-formaldehyde resins and unsaturated polyesters (OECD, 1994)
and in adhesives and coatings (WHO, 1994).
Assuming that the commercial octaBDE is not longer produced, the releases to the
environment must be associated to historical processes, as well as to releases during
14
the service life of articles containing the commercial mixtures and at the end of article
service life during disposal operations.
The information review by La Guardia et al (2006) allows estimations of the relative
contribution of each congener in different markets and time periods. As an example,
Figure 1 presents the calculations for European commercial products in 2001.
Relative contribution of PBDEs in European commercial formulas from 2001
1
0,1
0,01
0,001
0,0001
0,00001
BDE 17 BDE 28/33
BDE
47a/74
BDE 66/42 BDE 85
BDE 99
BDE 100
BDE 138
BDE 153
BDE 154
BDE
BDE 196 BDE 197
175/183a
BDE 206
BDE 207
BDE 209
Figure 1. Estimated relative contribution for the different BDE congeners in products in
the European market in 2001. Calculated from data published by La Guardia et al.,
2006. Note the logarithmic scale.
Although there are some figures on annual production of this mixture, there are no
accurate values on the amount of the commercial octa and/or the individual
homologues in articles in service and disposed at the world-wide level, but considering
the estimated figure of 6 000 tonnes/year (WHO, 1994) the total amount should be
expected in the 105 – 106 tonnes range. According to the BSEF, OctaBDE was
commercialized sometime in the mid 70’s. By the early 2000’s global production was
<4000 tonnes/year and by the time production ceased, demand was <500 tonnes.
While Thus, assuming 30 years of production at 6000 tonnes per year gives 180,000
tonnes, a figure within the proposed range.
In a 2002 document (Switzerland info) Switzerland reported for this country diffuse
emission from the use of products containing OctaBDE of about 0.37 t/a (based on
worst-case estimations) for a total stock of 680 tons.
2.2 Environmental fate
2.2.1 Persistence
No aerobic biodegradation of the hexa- to NonaBDEs is expected based on BIOWIN
estimates as recalcitrant with respect to biodegradation, and no degradation, based on
oxygen uptake, occurred in a 28-day closed bottle test (OECD 301D).
Gerecke et al. (2005) in a study on DecaBDE reported the degradation of nonaBDE
206 and 207 under anaerobic conditions using sewage sludge innoculum to OctaBDEs;
and this degradation has been confirmed in other studies (Gaul et al, 2006; He et al,
2006).
AOPWIN predicts half-lives for reaction with atmospheric hydroxyl radicals ranging
from 30.4 to 161.0 d for hexa- to NonaBDEs, respectively. In the atmosphere, octaBDE
15
is expected to strongly adsorb to suspended particles in the air and be removed via wet
and/or dry deposition. Note that predicted half-lives have not been empirically
substantiated, but are provided for reference purposes.
The photodecomposition of several BDEs has been studied in different matrices such
as methanol/water 80:20 (Eriksson et al. 2001) a sealed polyethylene tube exposed to
natural sunlight for up to 120 min (Peterman et al. 2003); or water (Sanchez-Prado et
al., 2006); in general degradation was faster for the higher brominated DEs than for the
lower brominated congeners. Rayne et al. (2006) suggest a short photochemical halflife for the hexa BDE153 in aquatic systems, with rapid photohydrodebromination to
some of the most prevalent penta- and tetra-brominated diphenyl ether congeners.
2.2.2 Bioaccumulation
Bioconcentration factors were reported by European Communities (2003) based on the
results of a study by CBC (1982), in which carp, Cyprinus carpio, were exposed for 8
weeks to commercial c-octaBDE at 10 or 100 µg/L using polyoxyethylene
hydrogenated castor oil as a dispersing agent. If it is assumed that the actual
concentrations of the c-octaBDE components were at or around the reported water
solubility for the substance of 0.5 µg/L, then the BCF for octaBDE would be <9.5 while
the BCF for heptaBDE would be about <1.1-3.8 and the BCF for c-octaBDE would be
about <10-36 (European Communities 2003). These BCF values are lower than would
be expected from the substance’s octanol-water partition coefficients. This was
potentially justified by a reduced bioavailability due to the inability of the large molecule
to cross cell membranes (European Communities 2003).
The UK has re-analyzed the CITI (1982b) bioconcentration data and suggests BCFs of
up to ~5,640 l/kg and ~ 2,580 l/kg for components D and E (both hexaBDPE).
However, toxicokinetic studies and monitoring data on humans and wildlife reviewed by
European Communities 2003, Canada Info 2 and others clearly demonstrate the
capability of the large BDE molecules to cross cell membranes. In fact UK info
indicates that studies on the levels of hexa- to octaBDE in the environment confirm the
presence of hepta and octaBDE isomers in some biota samples. Further data (see
below) confirms the bioavailability of large BDE molecules. Thus, the discussion on the
molecular size is useless and the evaluation should be related to the capability of BCFs
to quantify the bioaccumulation potential of these types of molecules (EU_SCHER,
2005).
In fact, oral exposure is expected to be the most relevant exposure pathway for these
chemicals. Van Beusekom et al. (2006) reported biota-sediment accumulation factors
between 1 and 3 for hexa and heptaBDE on two freshwater fish species in Spain and
concluded that 100% of the exposure was associated to food or food plus sediment for
bleak (Alburnus alburnus) and barbel (Barbus graellsii), respectively. The potential for
biomagnification has been demonstrated for hexa and heptaBDE (Burreau et al., 2004;
Sormo et al., 2006), and more recently suggested for the DecaBDE (Law et al., 2006).
The potential for bioaccumulation and biomagnification of these types of molecules can
be calculated using toxicokinetic models, based on metabolism and elimination.
Differences among isomers and the reported debromination processes introduce
additional uncertainty when reviewing field data.
16
Ciparis and Hale (2005) have reported a rapid bioaccumulation of hexaBDE in the
aquatic oligochaete, Lumbriculus variegates, exposed via sediment, with differences
between isomers and in the contamination pathway. A biota-sediment accumulation
factor of 9.1± 1.1 was observed for BDE 154, the highest concentration was found on
day 15 and the depuration rate constant was 0.032 ± 0.016 days-1.
Stapleton et al. (2004) in a dietary study on carps found depuration rates of 0.051±
0.036 days-1 and assimilation efficiencies of 4% ± 3 for the hexaBDE 153.
Stapleton and Baker (2003) and Stapleton et al. (2004b) in dietary studies on common
carp (Cyprinus carpio) found significant and rapid debromination of heptaBDE183 to
hexaBDE154 and to another unidentified hexaBDE congener within the intestinal
tissues of the carp after consuming its food. In vitro studies have demonstrated the
microsomal debromination in fish (Stapleton et al. (2006) and mammals (McKinney et
al., 2006).
The role of exposure levels in the elimination rate of several chemicals including
hexaBDE 153 has beeb study by the LPTC). Université Bordeaux I and the INIA’s
Laboratory for Ecotoxicology within the context of LRI-Cefic Research Project ECO1AINIA-1100. Depuration rates of 0.03-0.05 for Sparus aurata and Mytilus edulis, were
obtained (Alonso et al., 2006).
A recent study (Drouillard et al., 2007) has reported a depuration rate constant for the
hexaBDE 0.016 days-1 in juvenile American kestrels (Falco sparverius), with a
retention of about 50% of the administered dose.
A controlled feeding trial assessed transfer and accumulation of PBDEs from feed to
farmed Atlantic salmon (Salmo salar). On average, 95% of the total PBDE content in
the feed accumulated in whole salmon including heptaBDE 183 (Isosaari, et al. 2005).
2.2.3 Long range environmental transport
The presence of components of commercial octa BDE in remote areas (e.g. Norway
info, Norway Info 2; Canada info 2; Switzerland info2) is considered the best
demonstration for the potential for long range transport of these chemicals. As
debromination in the environment and biota has been suggested, hypothetically, the
presence of hexa to nonaBDEs could be explained by a long range transport of
decaBDE and its subsequent debromination, however, it is very unlikely to assume a
long range transport for decaBDE and not for the nona to hexa congeners.
Previous model predictions suggested a low potential for long-range atmospheric
transport for highly brominated BDEs (e.g. Wania and Dugani, 2004). However, in a
recent paper on DecaBDE, Breivik et al., (2006) have reported that chemicals that are
both sorbed to particles and potentially persistent in the atmosphere, such as BDE-209,
may have a larger potential for LRT than anticipated on the basis of earlier model
evaluations. This explanation could be also applied to c-OctaBDE components.
Recently Wegmann, et al (2007) applied the OECD Pov and LRTP Screening Tool to
the current POPs candidates, including c-octaBDE. The authors noted that they
believed that the substance property values for c-octaBDE in Wania and Dugani (2003)
were more accurate than the values in the POPRC document and therefore included
the Wania and Dugani values in their Monte Carlo uncertainty analysis. Although there
were considerable uncertainties, the results indicated that c-octaBDE has Pov and
LRTP properties similar to those of several known POPs.
17
2.3 Exposure

Summary of relevant information concerning exposure in local areas (both near
the source and in remote areas)
2.3.1 Atmosphere
Little information is available about concentrations of c-OctaBDE in the atmosphere. A
concentration of 52 000 pg/m3 was predicted for c-OctaBDE in the local atmosphere
resulting from emissions from polymer processing (EUSES predictions in European
Communities 2003).
Some measurements are available for PBDE congeners present in c-OctaBDE.
Strandberg et al. (2001) analyzed air samples from urban, rural and remote sites in the
United States near the Great Lakes. The average total c-OctaBDE-related congeners
(i.e., sum of BDEs 153, 154 and 190) present in the samples ranged from
approximately 0.2 to 0.9 pg/m3.
PBDEs (ranging from tri- to OctaBDEs) were detected in deposition samples collected
from sites in The Netherlands, Germany and Belgium, confirming their presence in
precipitation (Peters 2003). The PBDE composition of the samples could be linked to
the commercial penta- and OctaBDE mixes, with BDEs 47, 99 and 154 the
predominant congeners.
Bergander et al. (1995) analyzed air samples from two areas of Sweden remote from
industry for the presence of c-OctaBDE. No OctaBDE was detected in either the
particulate or gas phase samples (the detection limit not stated), but indications of the
presence of hexaBDE and heptaBDE were found in the particulate phase samples.
2.3.2 Water
Luckey et al. (2002) measured total PBDE (mono- to heptaBDE congeners)
concentrations of approximately 6 pg/L in Lake Ontario surface waters in 1999, with
hexaBDE congeners BDE153 and BDE154 each contributing approximately 5 to 8% of
the total.
C-OctaBDE was not detected in 1987 in 75 surface water samples taken in Japan at a
detection limit of 0.1µg/L or in 1988 in 147 water samples at a detection limit of 0.07
µg/L (Environment Agency Japan 1991). According to European Communities (2003),
the concentrations are considered to be representative of industrial, urban and rural
areas of Japan, but it is not known whether any of the sampling sites were in the
vicinity of a polybrominated diphenyl ether production site or a polymer processing site.
2.3.3 Sediments
Concentrations of c-OctaBDE in UK sediments ranged from <0.44 to 3030 µg/kg dw
(Allchin et al. 1999; Law et al. 1996). The highest levels were in sediments downstream
from a warehouse where c-DecaBDE was stored (Environment Agency 1997). COctaBDE was detected in 3 of 51 sediment samples from Japan in 1987 at
concentrations from 8 to 21 µg/kg (detection limit 7 µg/kg; ww or dw not specified), and
in 3 of 135 samples collected in 1988 at concentrations of 15 to 22 µg/kg (detection
limit 5 µg/kg; ww or dw not specified) (Environment Agency Japan 1991).
18
Kolic et al. (2004) presented levels of PBDEs in sediments from tributaries flowing to
Lake Ontario, and area biosolids in southern Ontario. Total hexa- and heptaBDEs (i.e.,
BDE 138, 153, 154 and 183) measured in sediment samples taken from fourteen
tributary sites (only 6 sites were reported) ranged from approximately 0.5 to 4.0 µg/kg
dw.
2.3.4 Soil
Hassanin et al. (2004) determined PBDEs in undisturbed surface soils (0-5 cm) and
subsurface soils from remote/rural woodland and grassland sites on a latitudinal
transect through the United Kingdom and Norway. In total, 66 surface soils were
analyzed for 22 tri- to heptaBDEs. Concentrations of total PBDEs in the surface soils
ranged from 0.065 to 12.0 µg/kg dw. Median PBDE concentrations in the surface soils
ranged from 0.61 to 2.5 µg/kg dw, with BDEs 47, 99, 100, 153 and 154 dominating the
total concentrations. The median concentration of the sum of these five congeners
ranged from 0.44 to 1.8 µg/kg dw. The researchers noted that the congener patterns in
the European background soils closely matched that reported for the c-pentaBDE
mixture. Northward along the latitudinal transect, there was an increasing relative
contribution of BDE 47 and other lighter PBDEs in comparison to the heavier PBDEs
measured in the samples.
2.3.5 Waste Effluent and Biosolids
Kolic et al. (2004) presented levels of PBDEs in sediments from tributaries flowing to
Lake Ontario, and of biosolids from nearby wastewater treatment facilities in southern
Ontario. Total hexa- and heptaBDEs (i.e., BDEs 138, 153, 154 and 183) measured in
biosolids ranged from approximately 111 to 178 µg/kg dw.
La Guardia (2001) analyzed 11 sewage sludge samples before land application from
Canada and the United States and found that total hexa- to OctaBDE congener
concentrations ranged from 40 to 2080 µg/kg dw. Kolic et al. (2003) investigated PBDE
levels in sewage sludge from 12 sites in southern Ontario and found hexa- to OctaBDE
congener concentrations totaled 124 to 705 µg/kg dw. Hexa- to OctaBDE congeners
were not detected in manure samples, and were at very low levels in pulp mill biosolids
(up to approximately 3 µg/kg dw).
Martinez et al. (2006) have recently reported concentrations of sum of hexa to
nonaBDE in the range of 15.5 to 160 µg/kg dw in sludge from municipal wastewater
treatment facilities in Spain, and up to 268 µg/kg dw in industrial facilities.
Gevao et al. (2006) measured PBDEs in coastal sediments receiving industrial and
municipal effluents in Kuwait. Total concentrations varied from 80 to 3800 pg/g dw with
heptaBDE183 dominating the congener distribution which resembled the commercial
formulation, Bromkal 79-8DE. Wastewater discharge from industrial activities appeared
to be the primary source of the compounds.
2.3.6 Biota
Concentrations of components found in c-OctaBDEs in biota were reviewed in Law et
al. (2003). The concentration of c-OctaBDE (reported as the commercial mixture DE79) in various biota found in aquatic environments in the UK ranged up to 325 µg/kg
ww in the liver of dab (Allchin et al. 1999). Concentrations of OctaBDE in muscle tissue
from UK fish ranged from <1 to 12 µg/kg ww (Allchin et al. 1999). In Japan, OctaBDE
19
was not detected in 75 fish samples taken in 1987 (detection limit 5 µg/kg ww), nor was
it detected in 144 fish samples taken from 48 locations in 1988-89 (detection limit 4
µg/kg; ww or dw not specified) (Environment Agency Japan 1991). HeptaBDE, along
with other PBDE congeners, was detected in eggs of peregrine falcons, Falco
peregrinus, from Sweden, at concentrations from 56 to 1300 µg/kg lipid (Lindberg et al.
2004).
Alaee et al. (1999) sampled lake trout from Lakes Superior, Huron and Ontario and
found that the total of hexaBDE and heptaBDE congeners ranged from an estimated
11 to 53 µg/kg lipid.
Rice et al. (2002) compared PBDE levels and congener patterns in carp and bass
sampled from two industrialized regions in the eastern U.S. The fish were collected
from the Detroit River, MI. and the Des Plaines River, IL. in May and June of 1999, and
analyzed for the presence of BDEs 47, 99, 100, 153, 154, 181, 183 and 190. Both river
systems are considered to receive high contributions from municipal and industrial
effluents. BDE47 dominated in fish taken from the Detroit River, comprising an average
of 53 to 56% of the total PBDEs by wet weight. BDEs 99, 100, 153 and 154 each
contributed between 8 and 9%, and BDEs 181 and 183 each comprised about 5% of
the total PBDEs. BDE190 was not detected in either fish species. Only carp were
sampled from the Des Plaines River, and these exhibited a markedly different PBDE
profile from that seen in the Detroit River fish. HeptaBDEs 181 and 183 were
predominant, contributing about 21% and 19%, respectively. BDE47 was third in
prevalence, comprising about 17% of the total PBDEs. Levels of the two hexaBDE
congeners, BDEs 153 and 154 were 8 to 13%, compared with about 5% for each of the
penta- congeners, BDEs 99 and 100. BDE190, not detected in the Detroit River fish,
was present at about 12% of total PBDE.
The congener profile identified in the Detroit River fish, with predominance of the tetraand pentaBDE congeners, was consistent with patterns reported in biota from other
parts of North America and the world. The greater prevalence of higher brominated
congeners evident in the Des Plaines River fish, however, was atypical. The authors
postulated that the unusual congener pattern displayed in fish from the Des Plaines
River may relate to the nature of wastewater discharges from manufacturing or waste
facilities in the region. The higher quantities of hexa- and heptaBDEs evident in the fish
samples may reflect higher discharge volumes of commercial OctaBDE products, so
that levels measured in fish represent a combination of commercial pentaBDE and
OctaBDE sources. The researchers note that the possible sources for the other
heptaBDEs, BDE 181 and BDE 190 that were found in the carp in Des Plaines River
are not obvious especially since no commercial products have been documented as
containing major quantities of these congeners. The authors speculate that the
significant presence of heptaBDE in the Des Plaines River fish may result from active
metabolism of BDE209 present in the river sediment; however river sediment
concentrations were not obtained in this study. They also suggest that differing
contributions to the two river systems from municipal wastewater treatment facilities
potentially played a role, but that congener determinations in effluent sources were also
not determined in this study.
Norstrom et al. (2002) evaluated the geographical distribution and temporal trends
(during the 1981 to 2000 period) of PBDEs in herring gull (Larus aargentatus) eggs
from a network of colonies scattered throughout the Great Lakes and their connecting
channels in 2000 (see Section 2.1.6.6 and Appendix D). Although samples were
analyzed for octa- to DecaBDE, these were not found at their respective limits of
detection (0.01-0.05 µg/kg ww). However, total concentrations of hexa- and heptaBDE
congeners (i.e., BDEs 153,154 and 183) increased 6 to 30 fold over the 1981 to 2000
20
period at the Lake Michigan (from 6.7 to 195.6 µg/kg ww), Lake Huron (from 13.8 to
87.6 µg/kg ww) and Lake Ontario (3.8 to 112.1 µg/kg ww) sites. This increase was not
as dramatic as that found for the tetra- and pentaBDE congeners.
Wakeford et al. (2002) conducted sampling of wild bird eggs in western and northern
Canada between 1983 and 2000. They determined that the total of hexa- and
heptaBDE congeners ranged from 0.148 to 52.9 µg/kg ww in Great Blue Heron (Ardea
herodias) eggs (on Canada’s west coast), 0.03 to 0.68 µg/kg ww in Northern Fulmer
(Fulmarus glacialis) eggs (in the Canadian arctic) and 0.009 to 0.499 µg/kg ww in Thick
Billed Murre (Uria lomvia) eggs (in the Canadian arctic). OctaBDE, nonaBDE and
DecaBDE congeners were subject to analysis by the researchers, but were not
detected (detection limit was not specified) in the any of the samples.
2.3.7 Humans
European Communities (2003) presents some information on the levels of components
of c-octaBDE measured in human samples. Large variations among individuals were
generally observed, but significant differences between the control population and
occupationally exposed groups were also reported.
In a recent study (Toms et al., 2007) the concentrations of PBDEs found in Australian
human milk were lower than those reported from North America but higher than those
reported from Europe and Asia

Summary of relevant information concerning exposure as a result of LRET
Measured levels of components of c-OctaBDE in biota from remote areas seem to be
the best available information for estimating exposure as result of LRET for these
chemicals. Knudsen et al (2005; Norway info) have recently review temporal trends of
PBDE in eggs from three bird species, three locations and three sampling times (from
1983 to 2003) from Northern Norway. Spatial differences were only observed for
hexaBDE 153, and increases in the measured concentration from 1983 to 2003 were
observed for the hexaBDE 153 and 154 and the heptaBDE 183. Mean values were
around 1 µg/kg ww for each isomer and maximum values above 10 µg/kg ww were
observed for BDE 154 and 183. Inter species differences could be associated to
feeding behavior and migration. In general the concentrations were lower than those
reported for similar species in industrialized areas and those observed in terrestrial
predatory birds.
Exposure to components of c-OctaBDE in remote areas is confirmed and based on the
available information should be attributed to a combination of releases and transport of
c-OctaBDE, c-pentaBDE (for hexaBDE) and c-DecaBDE (for nonaBDE), and to the
debromination of DecaBDE in the environment and biota. There is no sufficient
information for assessing these processes in quantified terms. The exposure route is
mainly via food, and even for water column animals water exposure is of low, if any,
relevance; therefore the BCFs are not suitable parameters for estimating the
bioaccumulation potential.
In addition to the feeding strategy, several additional confounding factors are
associated to the species to specific differences observed in the isomer distribution
pattern of PBDE in wildlife. These factors include, among others, species-specific
differences in assimilation, metabolism and depuration of different isomers, even with
the same level of bromination.
21
The presence of hexa and heptaBDE in fish from remote alpine lakes in Switzerland
(Switzerland info2) reported to be related to atmospheric deposition confirms the
potential for atmospheric long-range transport.

Information on bioavailability
Despite its large molecular size, the evidence demonstrates the capability of cOctaBDE components to cross the cellular membranes and to accumulate in biota.
Exposure from water is not relevant and significant assimilation rates have been
observed for oral and sediment exposures. Although the information is limited, the
assimilation and metabolisms of each isomer may vary significantly among species, but
also in relation to the administered dose. As a consequence, it is essential to
understand the toxicokinetics of these chemicals at environmentally relevant
concentrations.
These differences would justify the disparities observed in the assessment of
biomagnification potential for different trophic chains.
Like for other chemicals with similar properties, aging processes are expected to
reduce the bioavailability, and the experiments conducted on sediment dwelling
organisms comparing the bioaccumulation in spiked sediments and from contaminated
biosolids offer and indirect support for this hypothesis.
2.4 Hazard assessment for endpoints of concern
Experimental studies
Aquatic Organisms
The EU Risk Assessment report (European Communities 2003), presents a set of
studies on the commercial mixture and concludes that for water it seems sensible to
assume that no adverse effects on aquatic organisms are likely to occur at
concentrations up to the substance’s water solubility. However it must be noted, first,
that aquatic organisms are also exposed from food and/or sediment; and second, that
setting this strong conclusion on chemicals such as PBDEs requires multigenerational
or at least full life-cycle assays on the three taxonomic groups covering a large list of
sublethal effects, information which is unavailable at this time.
Benthic Organisms
There are two available 28 day spiked sediment studies on Lumbriculus variegatus
using the c-OctaBDE product (Great Lakes Chemical Corporation 2001a, b). These
studies found no statistically significant effects relevant to survival, reproduction or
growth at the highest tested concentration (1272 mg/kg dw and 1340 mg/kg dw
measured for sediments with 2.4% and 5.9% OC, respectively). Kinetic data from
Ciparis and Hale (2005) confirms the expected exposure and bioaccumulation under
these conditions.
Soil Organisms
Survival and growth of earthworms, Eisenia fetida, were not affected by a 56 day
exposure to a commercial OctaBDE formulation in an artificial soil at concentrations up
to 1470 mg/kg dw (measured concentration in sediments with 4.7% OC) (Great Lakes
Chemical Corporation 2001c).
22
The toxicity of c-OctaBDE to corn (Zea mays), onion (Allium cepa), ryegrass (Lolium
perenne), cucumber (Cucumis sativa), soybean (Glycine max), and tomato
(Lycopersicon esculentum) was evaluated in a 21-day emergence and growth study
using an artificial sandy loam soil (Great Lakes Chemical Corporation 2001d). No
statistically significant effects were observed for any plant species between the controls
and the treatments for emergence, survival or growth at any of the tested
concentrations (up to 1190 mg/kg dw, measured concentration).
Mammals and Birds
The lowest reported NOAEL for traditional endpoints is a NOAEL of 2 mg/kg/d based
on slight fetotoxicity at 5 mg/kg/d (considered relevant in the EU report) or 5 mg/kg
bw/d based on increased liver weights and decreased body weight gain among the
maternal treatment group and delayed fetal skeletal ossification at 15 mg/kg bw/d (for
those reviewers that do not consider relevant the slight fetotoxicity effects ) described
by Breslin et al. (1989) in a developmental toxicity study with Saytex 111 on New
Zealand White rabbits exposed orally via gavage over days 7 to 19 of gestation.
Effects on other endpoints have been described at lower concentrations, including:

A significant increase in EPN detoxification and p-nitroanEROD and isole
demethylation in male Sprague-Dawley rats at an oral dose of 0.60 mg/kg
bw/day OBDE formulation for 14-days.
 dose-dependent depletion of serum total thyroxine T4 and induced
pentoxyresorufin O-deethylase (PROD) activities in rats receiving 10 or more
mg/kg bw/day of commercial octabromo (Zhou et al. 2001)
Developmental neurotoxic effects. [COMMENT: Perhaps “developmental neurotoxic
effects” instead? This study is not adequately summarized here. This study was
conducted in male NMRI neonatal mice only. It is not entirely clear how many males
per dose group were exposed. There appeared to be around 19-24 animals per dose
group evaluated for the swim maze performances, but it was not clear how many were
evaluated for the other behavorial tests. Male mice were exposed by oral gavage on a
single day only, postnatal day 10, to 0, 0.45, 0.9, or 9.0 mg BDE 153 (hexaBDE) per kg
of body weight. The animals were then observed for spontaneous behavior
(locomotion, rearing, and total activity) at 2-, 4-, and 6-months of age, and the Morris
water maze test at 6-months of age. Measurement of nicotinic binding cites were also
evaluated in the hippocampus one week after completion of the behavioral tests.
Changes in spontaneous behavior (hyperactivity), impairments in learning and
memory, and reduced amounts of nicotinic receptors were observed and appeared to
get worse with age. While this study is useful for qualitative purposes as an indicator of
a concern for developmental neurotoxicity and for possible insights into the mechanism
of action of BDEs, it would not be considered by USEPA for quantitative purposes due
to several deficiencies in study design (for example, single gender, single exposure,
and uncertain number of animals exposed, among other things). End comment ]

Neonatal mice exposed to a single dose of 0.45 mg BDE153/kg bw on
postnatal day 10 showed when tested at 2, 4 and 6 months of age altered motor
behavior. Spatial learning ability and memory function in the adult mice were
also affected Viberg et al. (2001a)
 Eriksson et al. 2002a confirmed neurotoxic effects (aberrant behavioral
responses) on developing male mice exposed to 0.45 to 9.0 mg/kg bw of
BDE153 on day 10 of development. The effects were comparable to those
observed for PCB153 leading the authors to speculate that interactive
neurotoxic action may be possible between the two compounds.
 These neurotoxic effects have also been observed after a single oral dose of
nonaBDE 206 or OctaBDE 203 administered on postnatal day 3 or 10 to, or
PBDE 183; with disturbances in spontaneous behavior, leading to disrupted
23



habituation and a hyperactive condition in adults at the age of 2 months. (Viberg
et al., 2006).
Immunomodulation effects in captive nestling American kestrels (Falco
sparverius) have been reported by Fernie et al. (2005). Eggs within each clutch,
divided by laying sequence, were injected with safflower oil or penta-BDE
congeners-47, -99, -100, and -153 dissolved in safflower oil (18.7 microg
PBDEs/egg). For 29 days, nestlings consumed the same PBDE mixture
(15.6+/-0.3 ng/g body weight per day), reaching PBDE body burden
concentrations that were 120x higher in the treatment birds (86.1+/-29.1 ng/g
ww) than controls (0.73+/-0.5 ng/g ww). PBDE-exposed birds had a greater
PHA response (T-cell-mediated immunity), which was negatively associated
with increasing BDE-47 concentrations, but a reduced antibody-mediated
response that was positively associated with increasing BDE-183
concentrations. There were also structural changes in the spleen (fewer
germinal centers), bursa (reduced apoptosis) and thymus (increased
macrophages), and negative associations between the spleen somatic index
and PBDEs, and the bursa somatic index and BDE-47. Immunomodulation from
PBDE exposure may be exacerbated in wild birds experiencing greater
environmental stresses.
Fernie et al., 2006 also reported for the same species and test conditions that
exposure did not affect hatching or fledging success. PBDE-exposed nestlings
were larger (weight, bones, feathers) as they gained weight more quickly and
ate more food, the latter in association with their PBDE body burdens. BDE-100
was most influential on nestling growth, being positively associated with size,
weight gain, and food consumption. Increasing concentrations of BDE-183 and
-153 were related to longer bones and BDE-99 to longer feathers. The larger
size of the PBDE-exposed birds may be detrimental to their bone structure and
have excessive energetic costs.
In vitro studies indicates that BDE (including the hexaBDE 153) affected
protein kinase C (PKC) and calcium homeostasis in cerebellar granule neuronal
cultures in a similar way to those of a structurally-related polychlorinated
biphenyl (PCB) (Kodavanti et al., 2005)
Monitoring data on effects
There are several scientific papers comparing population effects observed in the field
with measured concentrations of POP like chemicals, including hexa to nonaBDE in
individuals from different species.
Unfortunately, wild populations are co-exposed to a mixture of PBDEs as well as to
other related brominated and chlorinated persistent pollutants, and with the current
level of knowledge epidemiological investigations can just present associations but no
cause-effect relationships between the exposure/accumulation of the components of
the commercial OctaBDE mixtures and potential adverse effects observed in wildlife.
A similar situation is observed regarding human health data, and no studies offering
conclusive evidence on the hazards of hexa to nonaBDE for humans at
environmentally relevant exposure levels have been found.
24
3 SYNTHESIS OF THE INFORMATION
The evaluation of the specific risks of commercial OctaBDE is complex and uncertain
as the consequence of:
 the presence of its components in commercial penta- and DecaBDE,
 the additional transformation in the environment through debromination, in
particular the evidence suggesting a significant role of debromination of OctaBDE
or DecaBDE to other PBDE congeners in biota is highly relevant as food is
expected to be the main exposure route for these chemicals, although increases
the difficulties for quantitative assessments, and
 mostly, because the lack of a solid body of toxicological and ecotoxicological
information for the mixture and its components covering the long-term low level
exposure conditions and the sublethal endpoints considered relevant for
assessing the risk of a POP candidate.
In this risk profile, hexa to nonaBDE have been considered the relevant components in
c-OctaBDE. It should be noted that other BDEs are also found in commercial mixtures,
but those are expected to be covered by the c-Penta entry and if and when there is
Stockholm POPs activity on c-Deca . It should be noted that theoretically this represent
80 different congeners, while the available information focuses on less than ten
congeners and some mixtures.
The persistence of these PBDE in the environment is well documented. The only
relevant degradation pathways identified until now are photolysis, anaerobic
degradation and metabolism in biota, acting through debromination and producing
other BDE which may have higher toxicity and bioaccumulation potential.
The bioaccumulation potential of these highly brominated BDEs cannot be described
by the BCF as waterborne exposure is of low if any relevance. As bioaccumulation is
the result of assimilation efficiency, metabolism and elimination rate, a reduced
assimilation does not necessarily result in low bioaccumulation potential. In fact, if
metabolisms and elimination rates are very low, the reduced assimilation will result in
longer times for achieving the steady state conditions, but for species with long life
spans a significant bioaccumulation may be expected.
The bioaccumulation potential for sediment exposure and particularly for exposure via
food is well documented for some hexa to nonaBDE. There is also enough toxicokinetic
information demonstrating that elimination rates in some vertebrate and invertebrate
species are equivalent to those observed for other POPs, with values in the range of
0.01 to 0.5 days-1, equivalent to a half life of about 14 to 70 days assuming first order
kinetic; and therefore, low enough for supporting a justified concern on the
bioaccumulation potential of Hexa to NonaBDE. Monitoring programs measuring PBDE
concentrations in biota conducted in industrialized and remote areas confirm this
potential for bioaccumulation.
It should be noted that differences in both assimilation and metabolism, and therefore
in the overall bioaccumulation potential, have been observed not only among
homologues, but also between isomers with the same level of bromination. Interspecies differences have also been reported. These differences may explain the
discrepancies in terms of food chain biomagnification potential described in the
literature.
25
In summary, a bioaccumulation potential is confirmed at least for some isomers, as well
as biomagnification in some food chains. As debromination into other POP-like
chemicals is expected to be a relevant contribution to the dissipation of hexa to
nonaBDE, the absence of food-chain biomagnification for a specific congener on a
specific taxonomic group does not necessarily decrease the overall concern.
In fact, biota monitoring data in remote areas offer the best demonstration on the
potential for long range transport of c-OctaBDE components, in particular for Hexa and
HeptaBDE. Theoretically this presence could also be explained by the transport of
DecaBDE and its subsequent debromination. However, the comparative analysis of the
available information on the physical-chemical properties of the different PBDE
homologues indicates that debromination from DecaBDE might contribute to the
process but it is not realistic to assume that this explains the process without additional
transport from other congeners. Thus, based on the available information a long-range
transport is expected for the c-OctaBDE components, and the role of atmospheric
transport is confirmed at least for Hexa and HeptaBDE based on its detection in alpine
lakes.
Unfortunately, the available information on the toxicity and ecotoxicity of hexa to
nonaBDE is very limited and does not offer enough information for presenting sound
toxicological and ecotoxicological profiles for each isomer, mixtures of isomers and
commercial mixtures.
No relevant effects have been observed in aquatic, sediment and soil laboratory
studies. The uptake of BDEs at least for the sediment exposure is expected within the
time-frame of the experiment, based on toxicokinetic studies. However, this information
cannot be used to conclude that Hexa to NonaBDE are not toxic for these organisms.
In fact, the measured endpoints and the exposure conditions, employed in these
assays are clearly insufficient for a proper assessment of chemicals such as hexa to
nonaBDE. Ecotoxicity tests on these types of chemicals should cover if possible
several generations or at least a full life cycle, and the measured endpoints must
include sublethal effects associated to the accumulation and re-mobilization of the
PBDEs during critical periods of development and reproduction, as well as the
ecologically relevant consequences of metabolic changes. In addition, all
environmentally relevant exposure routes must be addressed. The available tests do
not fulfill these conditions, thus, although no toxicity was reported, no concluding
statements on the toxicity of hexa to OctaBDE congeners for aquatic, sediment and soil
dwelling organisms can be presented.
The available information on mammals and birds offer relevant information. The lowest
reported NOAEL for traditional endpoints is 2-5 mg/kg bw/d based on slight fetotoxicity
or increased liver weights and decreased body weight gain among the maternal
treatment group and delayed fetal skeletal ossification. These effects are relevant for
the health and the ecological assessment and therefore useful for assessing risks for
humans and wildlife. Nevertheless, the additional available information also creates
concerns on the capability of these traditional endpoints for assessing the toxicological
profile of hexa to nonaBDE in mammals and other vertebrates.
The metabolic effects, their relevance and they level of coverage by the endpoints
measured in the experimental toxicity test should be considered.
However, the immuno-toxicological effects and particularly the delayed neurotoxic
effects observed after a single dose require specific attention. Although a quantitative
evaluation of these effects in terms of its potential risk for human health and ecosystem
is not possible based on the current level of information, the reported observations
26
must be analyzed with care. Certainly, the doses at which the effect have been
observed are well above exposure levels in remote areas estimated from current
monitoring data for a single congener. However, the effects have been observed for
different congeners, and realistic environmental exposure occurs for a mixture of
PBDEs. There is not enough information for considering if these effects may be
additive or even more than additive in synergistic exposures. The margins between
effects observed in the lab and estimated oral exposure levels in the field (based on
monitoring data) are not so high when the different isomers/homologues are sum.
McDonald (2005) estimated a critical body burden for hexa BDE 153 of 2000 µg/kg lipid
based on the NOEL of 0.45 mg/kg reported by Viberg et al 2003 and gives a margin of
safety of 7 between this level and the 95 percentile of total PBDE levels in US human
populations. It should be noted that hexa BDE 153 concentrations close to this value
have been found in several species and geographic sites (see Canada info 2 for a
review) and total PBDE concentrations frequently exceed largely this threshold.
Three additional concerns must be mentioned in the risk profile of PBDEs:



First, the reported debromination of highly brominated BDEs in the environment
and biota suggests a potential for the formation of congeners with demonstrated
POP properties such as those included in the risk profile of c-pentaBDE.
Second, there is an increasing evidence suggesting similar toxicological profiles
and therefore, equivalent hazards and concerns, between PBDEs and PCBs,
although the mode of action seems to be better categorized by AhRindependent mechanisms, as PBDEs do bind but not activate the AhR-AhR
nuclear translocator protein-XRE complex (Peters et al., 2006) and appear
capable of up-regulating CYP2B and CYP3A in rats at doses similar to that for
non-dioxin-like PCB153 (Sanders et al., 2005). As the persistence,
bioaccumulation potential and long range transport of the c-octaBDE
components are well documented, the confirmation of an equivalent level of
hazard for these two groups should be sufficient for confirming a long-range
transport associated risk
Third, the potential for formation of polybrominated dibenzo-p-dioxins and
furans (See European Communities, 2003 for a general discussion), although
not considered in this risk profile, should also be taken into account.
4 CONCLUDING STATEMENT
The evaluation of the human and environmental risk of commercial OctaBDE
associated to its potential for long range transport is not an easy task as the
commercial product is a mixture of components with different properties and profiles,
which may also be released to the environment due to its presence as components of
other PBDE commercial products and also produced in the environment by
debromination of commercial decaBDE.
Although the production of c-OctaBDE has ceased in developed countries and there is
no information suggesting that the chemical is produced elsewhere; it must be noticed
that the product is still present and released from articles in use and during their
disposal. Model estimations and measured levels in sewage sludge suggest that
current emissions are still significant.
The persistence of the hexa to nonaBDE is well documented and the main route of
degradation is debromination forming other BDEs, also of concern. The potential for
27
certain components in c-OctaBDE to bioaccumulate and also for biomagnification in
some trophic chains is also sufficiently documented and confirmed by the good
agreement between field observations in monitoring programmes and toxicokinetic
studies. Monitoring data in remote areas confirm the potential for long-range transport
and at least for some congeners the relevance of atmospheric distribution in this
process.
The highest difficulty appears for the estimation of the potential hazard of the
commercial mixture and its components. There are traditional ecotoxicological and
toxicological studies where no effects have been observed even at unrealistically high
concentrations. However, an in-depth assessment of these studies considering in
particular the properties and toxicokinetic of PBDE indicates that the test design,
exposure conditions and measured endpoints are not appropriate for a sound
assessment of these types of chemicals. Thus, the lack of effects reported in those
tests should be considered with care.
In addition, specific studies have reported particular hazards such as delayed
neurotoxicity and immunotoxicity which may be particularly relevant in the assessment
of both human health and ecosystem risks.
Based on the existing evidence, additional concerns related to the debromination into
toxic BDEs, the increasing evidence relating these chemicals with other POPs
(similarities between PBDEs and PCBs; relationships with dioxins and furans), and that
under Article 8, paragraph 7(a) of the Convention the lack of full scientific certainty shall
not prevent a proposal from proceeding, it is concluded that the components of cOctaBDE, Hexa to NonaBDE, are likely, as a result of LRET, to lead to significant
adverse human health and/or environmental effects, such that global action is
warranted.
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